EMEP/EEA air pollutant emission inventory guidebook

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1 Category Title NFR 5.C.1.a Municipal waste incineration SNAP Incineration of domestic or municipal wastes (without energy recovery) ISIC Version Guidebook 2016 Coordinator Carlo Trozzi Contributing authors (including to earlier versions of this chapter) Ole-Kenneth Nielsen, Malene Nielsen, Katja Hjelgaard, Peter Coleman, Otto Rentz, Dagmar Oertel, Haydn Jones, Michael Wenborn and Mike Woodfield EMEP/EEA air pollutant emission inventory guidebook

2 Contents 1 Overview Description of sources Process description Techniques Emissions Controls Methods Choice of method Tier 1 default approach Tier 2 technology-specific approach Tier 3 Emission modelling and use of facility data Data quality Completeness Avoiding double counting with other sectors Verification Developing a consistent time series and recalculation Uncertainty assessment Inventory quality assurance/quality control QA/QC Gridding Reporting and documentation Glossary References Point of enquiry EMEP/EEA air pollutant emission inventory guidebook

3 1 Overview This section includes the volume reduction, by combustion, of domestic and commercial refuse (often referred to as municipal solid waste (MSW)). Principally, this section includes the emissions from chimneys and duct work because of the availability of measurement data. Care must be taken to prevent double counting of emissions reported here and in the relevant combustion chapter in the relevant source category in 1.A. All the activities and emission factors with regard to the incineration of waste are explained in the waste incineration chapters. If there is heat recovery in the incineration process, it is good practice to report the emissions in the relevant combustion sector in 1.A. If no heat recovery is applied, it is good practice to report the emissions under the appropriate waste incineration sector. The emissions of compounds such as volatile organic compounds (VOCs), sulphur dioxide, hydrogen chloride and particulate matter (PM) from waste incineration are unlikely to contribute significantly to total emissions. However, waste incinerators have been a major source of emissions of polychlorinated dibenzo-dioxins and polychlorinated dibenzo-furans PCDD/Fs, other persistent organic pollutants (POPs) and some heavy metals such as cadmium and mercury (Leech, 1993). MSW incinerators in many countries now apply extensive abatement techniques and comply with emission limits, and in these cases the contribution of MSW incinerators to total emissions of PCDD/Fs and heavy metals has greatly decreased. 2 Description of sources 2.1 Process description Municipal solid waste is the unwanted material collected from households and commercial organisations. It consists of a mix of combustible and non-combustible materials, such as paper, plastics, food waste, glass, defunct household appliances and other non-hazardous materials. The quantity produced per person varies with the effectiveness of the material recovery scheme in place and with the affluence of the neighbourhood from which it is collected. Municipal waste can be incinerated to: reduce its volume; save landfill space and costs; recover energy from its combustion, either for district/process heating and/or for electricity generation. Figure 2-1 shows a process scheme for the incineration of municipal waste. Only combustion emissions arise from the incinerator. It is good practice to report the emissions accordingly: in the relevant combustion source category when energy recovery is applied (when the incinerated waste is used as a fuel for another combustion process); in this source category when no energy recovery is applied. EMEP/EEA air pollutant emission inventory guidebook

4 Fuel 5.C.1.a Municipal waste incineration Figure 2-1 Process scheme for source category 5.C.1.a Municipal waste incineration, with energy recovery (left panel) and without energy recovery (right panel) Incinerator Waste Incinerator 2.2 Techniques There are many different furnace designs and combustion techniques in use in Europe for MSW incineration. However, the main influences on the total emission expected from these incinerators are the waste burning capacity of the incinerator, the type of incinerator (mass burn excess air or modular starved air), the way in which it is operated (e.g. whether it includes heat recovery) and the degree of abatement fitted to the plant. Figure 2-2 shows a simple diagram of the components of a typical MSW incinerator. EMEP/EEA air pollutant emission inventory guidebook

5 Figure 2-2 Components of a typical mass burn, excess air MSW incinerator Secondary air Secondary combustion chamber (radiant shaft) Further heat recovery (convection boiler) Crane Feed hopper Heat recovery Stack Waste Primary air Grate Gas cleaning There are 3 key classes of MSW incineration technology which depend on the quantity and form of the waste burned. These are mass burn units, modular combustors and fluidised bed combustors. Mass burn units In mass burn units, the MSW is incinerated without any pre-processing other than the removal of items too large to go through the feed system and removal of hazardous items, e.g. compressed gas cylinders. Mass burn combustors usually range in size from e.g. 45 to 900 tonnes waste/day. Operation of mass burn units typically includes the introduction of excess air. Designs of mass burn combustors include mass burn water wall, mass burn rotary water wall combustor, and mass burn refractory wall. Modular combustors Modular combustors are similar to mass burn combustors as they burn waste that has not been preprocessed, but they are typically shop fabricated and generally smaller, ranging in size from 4 to 130 tonnes waste/day. One of the most common types of modular combustors is the starved air or controlled air type. They are used where start-ups occur each day and/or where throughputs are low, for example at commercial/factory sites or in rural areas. Fluidised bed combustors (FBC) Fluidised bed combustors have a bed of sand or similar inert material which is agitated or fluidised by an upward flow of air through a porous plate below it. Combustion occurs within the bed. For the combustion of MSW in FBC, the fuel has to be treated (e.g. shredded) in order to obtain a suitable size. Waste, in whatever form, enters the combustion chamber via the feeder hopper. In a typical incinerator, refuse is placed on a grate that moves the waste through the combustor, mixing the waste thoroughly with the hot air to ensure effective combustion. Grate-firing installations are capable of burning a range of wastes, which is useful as the composition of the waste varies widely. They can also operate at a range of flow rates. Apart from fluidised bed, there are two main types of grate: moving grate; rotary furnace. EMEP/EEA air pollutant emission inventory guidebook

6 The main combustion technique used for the incineration of MSW is the moving grate. Fluidised bed combustion (FBC) or rotary furnace techniques have had a more limited use for the incineration of MSW. Many incinerator designs have two combustion chambers. Air is supplied to the primary chamber through the waste (primary air). The incomplete combustion products (CO and organic compounds) pass into the secondary combustion chamber where additional air (secondary air) is added and combustion is completed. Incinerator size Small incinerator plants with a restricted waste supply are often operated as batch processes. This increases the frequency of start up and burn out emissions which are often excessive. 2.3 Emissions As well as persistent organic pollutants (e.g. dioxins), and some heavy metals (e.g. Pb, Cu, Cd, Cr, Ni, Hg), pollutants released are sulphur oxides (SOx), nitrogen oxides (NOx), volatile organic compounds (non-methane VOCs), carbon monoxide (CO) and ammonia (NH3). Carbon monoxide emissions result when carbon in the waste is not oxidised to carbon dioxide (CO2). High levels of CO indicate that the combustion gases were not held at a sufficiently high temperature in the presence of oxygen (O2) for a long enough time to convert CO to CO2. Because O2 levels and air distributions vary among combustor types, CO levels also vary among combustor types. Carbon monoxide concentration is a good indicator of combustion efficiency, and is an important criterion for indicating instabilities and non-uniformities in the combustion process (US Environmental Protection Agency (US EPA), 1995). Nitrogen oxides are products of all fuel/air combustion processes. Nitric oxide (NO) is the primary component of NOx; however, nitrogen dioxide (NO2) and nitrous oxide (N2O) are also formed in smaller amounts. Nitrogen oxides are formed during combustion through oxidation of nitrogen in the waste, and oxidation of atmospheric nitrogen. Conversion of nitrogen in the waste occurs at relatively low temperatures (less than C), while oxidation of atmospheric nitrogen occurs at higher temperatures. Because of the relatively low temperatures at which municipal waste furnaces operate, 70 to 80 percent of NOx formed in municipal waste furnaces is associated with nitrogen in the waste. A variety of organic compounds, including chlorobenzenes, polychlorinated biphenyls (PCB), polycyclic aromatic hydrocarbons (PAH) and PCDD/Fs are present in MSW or can be formed during the combustion and post-combination processes. Organics in the flue gas can exist in the vapour phase or can be condensed or absorbed on fine particulates. 2.4 Controls The level of abatement at an incinerator plant varies, depending on the size of the plant, emission regulations, etc. Modern plants, and many older plants which have been updated, have a range of different emission abatement equipment which aim to ensure compliance with emission regulations and address the three main environmental impacts of waste incineration: acid gas, heavy metal and dioxin emissions. Typical approaches used include: fabric filters (particle control); electrostatic precipitators (particle control); EMEP/EEA air pollutant emission inventory guidebook

7 wet scrubbers (acid gas removal); semi-dry scrubbers/spray absorber systems (acid gas removal); dry injection systems (acid gas removal); adsorption using activated carbon/activated lignite coke (PCDD/F and mercury removal). These control systems are described in the glossary. They are commonly needed in combination; the fabric filter has a secondary function for acid gas control and similarly the wet scrubber for particle control. NOx emissions are controlled by using primary or secondary measures as described in chapter 1.A.1.a, Public electricity and heat production (Combustion in energy and transformation industries chapter). In the past, many small incinerators have had negligible emission control equipment and the older large plants have had particle control only, frequently by electrostatic precipitator. This abates emissions of heavy metals but may increase the PCDD/F emissions over unabated plant. Older plants also have less ash burn out as the waste combustion is less efficient and this reduces the carbon dioxide emission factor. Although later decay of the ash may lead to carbon dioxide and VOC emission, this has not been considered here. Today, more comprehensive abatement techniques have become common as many countries must now apply with legislation such as the EU waste incineration directive. 3 Methods 3.1 Choice of method Figure 3-1 presents the procedure to select the methods for estimating emissions from incineration of industrial wastes. The basic idea is: if detailed information is available, use it; if the source category is a key category, a Tier 2 or better method must be applied and detailed input data must be collected. The decision tree directs the user in such cases to the Tier 2 method, since it is expected that it is more easy to obtain the necessary input data for this approach than to collect facility level data needed for a Tier 3 estimate; the alternative of applying a Tier 3 method, using detailed process modelling, is not explicitly included in this decision tree. However, detailed modelling will always be done at facility level and results of such modelling could be seen as facility data in the decision tree. EMEP/EEA air pollutant emission inventory guidebook

8 Figure 3-1 Decision tree for source category 5.C.1.a Municipal waste incineration Start Facility data Available? Yes All incineration covered Yes Use Tier 3 Facility data only No No Use Tier 3 Facility data & extrapolation Technology Stratification available? Yes Use Tier 2 technology specific activity data and EFs No Key source? Yes Get technology stratified activity data and EFs No Apply Tier 1 default EFs 3.2 Tier 1 default approach Algorithm The simpler methodology relies on the use of a single emission factor for each pollutant species, combined with a national waste incineration statistic. The general equation can be written as: E pollutant AR EF (1) production pollutant This equation is applied at the national level. Information on the production statistics can be obtained from the national annual quantity of municipal waste incinerated. The Tier 1 emission factors assume an averaged or typical technology and abatement implementation in the country. In cases where specific abatement options are to be taken into account, a Tier 1 method is not applicable and a Tier 2 or Tier 3 approach must be used Default emission factors Table 3-1 presents the Tier 1 default emission factors for the incineration of municipal wastes. For the Tier 1 emission factors, it is assumed that desulphurisation, NOx abatement (SNCR), particle abatement (ESP and/or FB) and activated carbon are in place. These emission factors can be assumed to be representative for modern waste incineration plants and are based on measurements carried out in EMEP/EEA air pollutant emission inventory guidebook

9 Denmark (Nielsen et al., 2010) following the implementation of the EU waste incineration directive. The original emission factors are based on energy input and have been converted using a net calorific value (NCV) of 10.5 GJ per tonnes. 95 % confidence intervals are estimated by expert judgement. Table 3-1 Tier 1 emission factors for source category 5.C.1.a Municipal waste incineration Tier 1 default emission factors Code Name NFR source category 5.C.1.a Municipal waste incineration Fuel NA Not applicable Not estimated Pollutant Value Unit 95 % confidence interval Reference Lower Upper NO x 1071 g/mg Nielsen et al. (2010) CO 41 g/mg Nielsen et al. (2010) NMVOC 5.9 g/mg Nielsen et al. (2010) SO 2 87 g/mg Nielsen et al. (2010) NH g/mg Nielsen et al. (2010) TSP 3.0 g/mg Nielsen et al. (2010) PM g/mg CEPMEIP PM g/mg CEPMEIP BC % of PM Olmez et al. (1988) Pb 58.0 mg/mg Nielsen et al. (2010) Cd 4.6 mg/mg Nielsen et al. (2010) Hg 18.8 mg/mg Nielsen et al. (2010) As 6.2 mg/mg Nielsen et al. (2010) Cr 16.4 mg/mg Nielsen et al. (2010) Cu 13.7 mg/mg Nielsen et al. (2010) Ni 21.6 mg/mg Nielsen et al. (2010) Se 11.7 mg/mg Nielsen et al. (2010) Zn 24.5 mg/mg Nielsen et al. (2010) PCBs 3.4 ng/mg Nielsen et al. (2010) PCDD/F 52.5 ng/mg Nielsen et al. (2010) Benzo(a)pyrene 8.4 µg/mg Nielsen et al. (2010) Benzo(b)fluoranthene 17.9 µg/mg Nielsen et al. (2010) Benzo(k)fluoranthene 9.5 µg/mg Nielsen et al. (2010) Indeno(1,2,3-cd)pyrene 11.6 µg/mg Nielsen et al. (2010) HCB 45.2 µg/mg Nielsen et al. (2010) Activity data For the simpler methodology the national annual incineration of waste is required. In addition, a more reliable estimate can be made if information is available on the typical levels of abatement technology used and on the associated overall abatement efficiency. Emission factors are presented in mass per unit mass of waste burned. For recalculation in terms of energy (g/gj), a default NCV (net calorific value) is available from the Introduction of the Energy volume of the 2006 Intergovernmental Panel on Climate Change (IPCC) Guidelines (IPCC, 2006) and is 10 TJ/Gg (range 7 18 TJ/Gg). ( 1 ) For the purposes of this guidance, BC emission factors are assumed to equal those for elemental carbon (EC). For further information please refer to Chapter 1.A.1 Energy Industries. EMEP/EEA air pollutant emission inventory guidebook

10 3.3 Tier 2 technology-specific approach Algorithm The Tier 2 approach is similar to the Tier 1 approach. To apply the Tier 2 approach, both the activity data and the emission factors need to be stratified according to the different techniques that may occur in the country. The approach followed to apply a Tier 2 approach is as follows. Stratify the waste incineration in the country to model the different product and process types occurring in the national waste incineration industry into the inventory by: defining the production using each of the separate product and/or process types (together called technologies in the formulae below) separately; and applying technology specific emission factors for each process type: E AR, EF (2) pollutant technologi es productiontechnology technology,pollutant where: ARproduction,technology = the production rate within the source category, using this specific technology, EFtechnology,pollutant = the emission factor for this technology and this pollutant. A country where only one technology is implemented will result in a penetration factor of 100 % and the algorithm reduces to: E pollutant AR EF (3) production technology,pollutant where: Epollutant = the emission of the specified pollutant, ARproduction = the activity rate for the waste incineration, EFpollutant = the emission factor for this pollutant. The emission factors in this approach still will include all sub-processes within the waste incineration. EMEP/EEA air pollutant emission inventory guidebook

11 3.3.2 Technology-specific emission factors The table below lists the uncontrolled emission factors for use with municipal or domestic waste incineration activities. The abatement efficiencies in subsection of the present chapter may be used to calculate appropriate emission factors when abatement is in place. Table 3-2 Tier 2 emission factors for source category 5.C.1.a Municipal waste incineration Tier 2 emission factors Code Name NFR Source Category 5.C.1.a Municipal waste incineration Fuel NA SNAP (if applicable) Incineration of domestic or municipal wastes (without energy recovery) Technologies/Practices Region or regional conditions Abatement technologies uncontrolled Not applicable Not estimated NH 3, Se, Indeno(1,2,3-cd)pyrene Pollutant Value Unit 95% confidence interval Reference Lower Upper NO x 1.8 kg/mg waste Guidebook (2006) CO 0.7 kg/mg waste Guidebook (2006) NMVOC 0.02 kg/mg waste Guidebook (2006) SO kg/mg waste Guidebook (2006) TSP 18.3 kg/mg waste Guidebook (2006) PM kg/mg waste Guidebook (2006) PM kg/mg waste Guidebook (2006) BC % of PM Olmez et al. (1988) Pb 104 g/mg waste Guidebook (2006) Cd 3.4 g/mg waste Guidebook (2006) Hg 2.8 g/mg waste Guidebook (2006) As 2.14 g/mg waste US EPA (1996) Cr g/mg waste Morselli et al. (2002) Cu g/mg waste Morselli et al. (2002) Ni 0.12 g/mg waste Morselli et al. (2002) Zn 0.9 g/mg waste Morselli et al. (2002) PCBs 5.3 mg/mg waste Guidebook (2006) PCDD/F 3.5 mg I-TEQ/Mg waste 2 7 UNEP (2005) Benzo(a)pyrene 4.2 mg/mg waste Guidebook (2006) Benzo(b)fluoranthene 3.2 mg/mg waste Guidebook (2006) Benzo(k)fluoranthene 3.1 mg/mg waste Guidebook (2006) HCB g/mg waste Berdowski et al. (1997) Note: The source of these numbers only lists the emission factor sum: benzo(bk)fluoranthene has an emission factor of 6.3 mg/mg municipal waste burned Abatement A number of add-on technologies exist that are aimed at reducing the emissions of specific pollutants. The resulting emission can be calculated by replacing the technology specific emission factor with an abated emission factor as given in the formula: EF technology, abated ( 1 abatement) EFtechnologyunabated, (4) This section presents default abatement efficiencies for a number of different abatement techniques applied in the municipal waste incineration. Additional information on PM and heavy metal emission ( 2 ) For the purposes of this guidance, BC emission factors are assumed to equal those for elemental carbon (EC). For further information please refer to Chapter 1.A.1 Energy Industries. EMEP/EEA air pollutant emission inventory guidebook

12 factors with abatement in place is available from US EPA AP42, Chapter 2, Section 1 on Refuse Combustion (US EPA, 1996). Most of the abatement efficiencies are derived from an assessment of abated emission factors in earlier versions of the Guidebook. No full literature references are provided. The abatement efficiencies of dioxins and furans (PCDD/F) with a description mentioning Air Pollution Control (APC) are taken from the United Nations Environment Programme (UNEP) Chemicals Toolkit for Dioxins and Furans (UNEP, 2005). These are related to a low technology combustion plant without APC system, which has a PCDD/F emission factor of μg TEQ/Mg MSW burned (see Tier 2 technologyspecific emission factor table). Table 3-3 Abatement efficiencies (ηabatement) for source category 5.C.1.a Municipal waste incineration Tier 2 Abatement efficiencies Code Name NFR Source Category 5.C.1.a Industrial waste incineration Fuel NA not applicable SNAP (if applicable) Incineration of industrial wastes Abatement technology Pollutant Efficiency 95% confidence interval Reference Default Value Lower Upper Acid gas abatement SO2 76% 29% 92% Guidebook (2006) Particle abatement only TSP 98% 95% 99% Guidebook (2006) PM10 98% 95% 99% Guidebook (2006) PM2.5 98% 95% 99% Guidebook (2006) Particle and acid gas abatement TSP 99.99% 99% 99.99% Guidebook (2006) PM % 99% 99.99% Guidebook (2006) PM2.5 99% 98% 99.99% Guidebook (2006) EU Waste Incineration Directive TSP 97% 91% 99% Guidebook (2006) (WID) compliant plant PM10 61% 0% 87% Guidebook (2006) PM2.5 99% 98% 99.99% Guidebook (2006) Controlled combustion; minimal PCDD/F 90% 70% 97% UNEP (2005) APC system Controlled combustion; good PCDD/F 99% 97% 99.99% UNEP (2005) APC system High technology combustion; sophisticated APC system PCDD/F 99.99% 99.99% 99.99% UNEP (2005) Note: WID compliant plant: half hourly limit concentration of 10 mg/m 3 at 11 % oxygen, from BAT reference document (European Commission, 2006) Activity data For industrial waste incineration, the national annual quantity of industrial waste incinerated is required. Subsequently, for sludge incineration, the national annual incineration of sewage sludge is required. Emission factors are presented in mass per unit mass of waste burned. For recalculation in terms of energy (g/gj), a default NCV (net calorific value) is available from the Introduction of the Energy volume of the 2006 IPCC Guidelines (IPCC, 2006) and is 10 TJ/Gg (range 7 18 TJ/Gg). 3.4 Tier 3 Emission modelling and use of facility data A Tier 3 method is not available for this source. EMEP/EEA air pollutant emission inventory guidebook

13 4 Data quality 4.1 Completeness Care should be taken to include emissions from waste incineration either in this source category, or in the relevant 1.A combustion chapter. It is good practice to check if this is indeed the case. 4.2 Avoiding double counting with other sectors Care should be taken not do double count emissions from waste incineration. It is good practice to check that emissions not included in this source category (because the heat from the incineration is recovered and the waste is subsequently used as a fuel) are reported in the relevant 1.A combustion chapter. 4.3 Verification Best Available Technique emission factors The IPPC Reference Document on Best Available Techniques on Waste Incineration (European Commission, 2006) describes achievable emission levels and the technologies necessary to achieve those levels in the process of waste incineration. However, no specific emission limit values for municipal waste incineration are given in this document. Some generic emission concentrations for waste incineration are given in the table below. More information is available from the BREF document for Best Available Techniques in Waste Incineration (European Commission, 2006). Table 4-1 BAT compliant emission factors for source category 5.C.1.a Municipal waste incineration BAT compliant emission factors Code Name NFR Source Category 5.C.1.a Municipal waste incineration Fuel NA not applicable 95% confidence interval Pollutant Value Unit Lower Upper SO mg/nm3 NO2 (using SCR) mg/nm3 NO2 (not using SCR) mg/nm3 CO 5-30 mg/nm3 Hg mg/nm3 PCDD/F mg I-TEQ/Nm3 TSP 1-5 mg/nm3 NH3 < 10 mg/nm3 4.4 Developing a consistent time series and recalculation No specific issues. 4.5 Uncertainty assessment It is good practice to consider that from country to country the composition of the incinerated waste may vary due to differences in waste definitions and fractionation. This could lead to country-specific emission factors that are not comparable to those of other countries. EMEP/EEA air pollutant emission inventory guidebook

14 4.5.1 Emission factor uncertainties Emission factors are likely to vary considerably between different incinerators, depending on the operating conditions and on which of the many combinations of gas cleaning equipment is in use on the plant. The variability at just a single plant for PCDD/Fs, for example, can be an order of magnitude between different sampling periods. The ranges in emission factors and the data quality ratings (mainly C, D or E) demonstrate the high uncertainty Activity data uncertainties No specific issues. 4.6 Inventory quality assurance/quality control QA/QC No specific issues. 4.7 Gridding No specific issues. 4.8 Reporting and documentation No specific issues. 5 Glossary Municipal solid waste (MSW) Mass burn units Mass burn water wall Mass burn rotary water wall Mass burn refractory Modular combustors Refuse-derived fuel (RDF) combustors Moving grate Fluidised bed combustors (FBC) Energy recovery PAHs PCBs PCDD/Fs A mix of unwanted waste material from households and commercial organisations. Incinerators which burn waste without any major pre-processing. These are typically fed with excess air. Designs have water-filled tubes in the furnace walls that are used to recover heat for production of steam and/or electricity. Combustors use a rotary combustion chamber constructed of water-filled tubes followed by a water wall furnace. Designs are older and typically do not include any heat recovery. Similar to mass burn units, but are generally pre-fabricated and smaller, and are typically starved air. Incinerate processed waste (e.g. waste that has been sorted, shredded, pelletized, etc.). A grate on which the waste is burned. Primary air is introduced through the grate and passes through the mass of waste material. The moving grate agitates the waste and promotes thorough distribution of air. Have a bed of sand or similar inert material which is agitated or fluidised by an upward flow of air through a porous plate below it. Combustion occurs within the bed. MSW is only burned if it has been sorted or shredded (i.e. as RDF). The removal of heat from the exhaust gases so as to provide heat and/or electricity for use in the plant or elsewhere. Polycyclic aromatic hydrocarbons. Polychlorinated biphenyls. Polychlorinated dibenzo-para-dioxins and polychlorinated dibenzo furans a series of chlorinated aromatic compounds, commonly known as dioxins. EMEP/EEA air pollutant emission inventory guidebook

15 POPs NMVOCs HCB Fabric filters/filter bags (FB) Electrostatic precipitators (ESP) Wet scrubbers Semi-dry scrubbers/ spray absorber systems (spray drying) Dry injection systems Adsorption using activated carbon/ activated lignite coke Persistent organic pollutants. Non-methane volatile organic compounds. Hexachlorobenzene. Consist of semi-permeable material in the form of bags or sleeves which trap particles and which are mounted in an airtight housing (baghouse) which is divided into a number of sections. Fabric filters are also used as a second stage in acid gas control systems. Use the principle of electrostatic attraction to remove entrained particles from the flue gases. They consist of rows of discharge electrodes (wires or thin metal rods), through which a high voltage is applied, and which run between an array of parallel rows of metal plates which collect the charged particles. Remove acid gases (e.g. HCl, HF and SO 2) by washing the flue gases in a reaction tower. Designed to provide a high gas-liquid contact. In the first stage the gases are cooled by water sprays, removing HCl, HF, some particulates and some heavy metals. In the second stage calcium hydroxide or another suitable alkali is used to remove SO 2 and any remaining HCl. Make use of an alkaline reagent slurry (usually calcium hydroxide) which is introduced as a spray of fine droplets. The acid gases are absorbed into the aqueous phase on the surface of these droplets and neutralised to form a dry product, which is collected in an electrostatic precipitator or fabric filter. Involve the injection of an alkaline reagent (e.g. calcium hydroxide or sodium bicarbonate) as a fine, dry powder to remove and neutralise acid gases. The neutralised product is normally collected in a fabric filter. Several different technologies have been developed for dioxin and mercury control. These systems can also be fairly effective at removing HCl and SO 2 and act as a useful polisher for these acid gases. EMEP/EEA air pollutant emission inventory guidebook

16 6 References Berdowski J.J.M., Baas J, Bloos JP.J., Visschedijk A.J.H., Zandveld P.Y.J. (1997). The European Atmospheric Emission Inventory for Heavy Metals and Persistent Organic Pollutants. Umweltforschungsplan des Bundesministers fur Umwelt, Naturschutz und Reaktorsicherheit. Luftreinhaltung. Forschungbericht /03. TNO, Apeldoorn, The Netherlands. CEPMEIP. The Coordinated European Particulate Matter Emission Inventory Programme (CEPMEIP) database. Netherlands Organisation for Applied Scientific Research (TNO). Data collected Available via European Commission (2006). Integrated Prevention and Pollution Control. Reference Document Best Available Techniques for waste incineration, August Guidebook (2006). European Monitoring and Evaluation Programme (EMEP)/Corinair Emission Inventory Guidebook, version 4 (2006 edition), published by the European Environmental Agency. Technical report No 11/2006. Available via IPCC (2006). Intergovernmental Panel on Climate Change Leech (1993). UK Atmospheric Emissions of Metals and Halides , Warren Spring Laboratory Report LR 923, Department of Trade and Industry, London UK. Morselli L., Passarini F. and Bartoli M. (2002). The environmental fate of heavy metals arising from a MSW incineration plant, Waste Management 22, pp Nielsen, M., Nielsen, O.-K. & Thomsen, M. 2010: Emissions from decentralised CHP plants Energinet.dk Environmental project no. 07/1882. Project report 5 Emission factors and emission inventory for decentralised CHP production. National Environmental Research Institute, Aarhus University. 113 pp. NERI Technical report No Available via Olmez, I., Sheffield, A.E., Gordon, G.E., Houck, J.E., Pritchett, L.C., Cooper, J.A., Dzubay T.G. & Bennett, R.L., 1988: Compositions of Particles from Selected Sources in Philadelphia for Receptor Modeling Applications. JAPCA 38: (1988). UNEP (2005). United Nations Environmental Programme, PCDD/PCDF Toolkit US EPA (1995). Compilation of Air Pollutant Emission Factors AP42 (CD-Rom). US EPA (1996). United States Environmental Protection Agency, AP42, fifth edition, Chapter 2, Section 1: Refuse Combustion. US EPA, Office of Air Quality Planning and Standards, Research Triangle Park, North Carolina. 7 Point of enquiry Enquiries concerning this chapter should be directed to the relevant leader(s) of the Task Force on Emission Inventories and Projection s expert panel on combustion and industry. Please refer to the TFEIP website ( for the contact details of the current expert panel leaders. EMEP/EEA air pollutant emission inventory guidebook